Comparison of Ten Metal-Doped LaFeO3 Samples on Photocatalytic Degradation of Antibiotics in Water under Visible Light: Role of Surface Area and Aqueous Phosphate Ions

Doping semiconducting oxides, such as LaFeO3 (LF), with metallic elements is a good strategy to improve the performance of photocatalysts. In this study, LF and ten different nanopowders metal-doped at the La or Fe site of LaFeO3 were evaluated in the photocatalytic degradation of ciprofloxacin (CP) and oxytetracycline (OTC). The following metals were used in the doping (mol%) process of LF: Pd 3% and 5%; Cu 10%; Mg 5%, 10%, and 20%; Ga 10%; Y 10% and 20%; and Sr 20%. The doped samples were synthetized using a citrate auto-combustion technique. From the X-ray diffraction (XRD) data, only a single crystalline phase, namely an orthorhombic perovskite structure, was observed except for trace amounts of PdO in the sample with Pd 5%. The specific surface area (SSA) ranged from 9 m2 g−1 (Ga 10%) to 20 m2 g−1 (Mg 20%). SEM images show that all samples were constituted from agglomerates of particles whose sizes ranged from ca. 20 nm (Mg 20%) to ca. 100 nm (Pd 5%). Dilute aqueous solutions (5 × 10−6 M) prepared for both CP and OTC were irradiated for 240 min under visible-light and in the presence of H2O2 (10−2 M). The results indicate a 78% removal of OTC with Cu 10% doped LF in a phosphate buffer (pH = 5.0). The degradation of CP is affected by pH and phosphate ions, with 78% (in unbuffered solution) and 54% (in phosphate buffer, pH = 5.0) removal achieved with Mg 10% doped LF. The reactions follow a pseudo-first order kinetic. Overall, this study is expected to deepen the assessment of photocatalytic activity by using substrates with different absorption capacities on photocatalysts.


Introduction
Besides conventional wastewater treatment methods, the application of advanced oxidation processes (AOPs) has received widespread attention for decades. AOPs are based on the formation and reaction of reactive oxidation species (ROS), mostly generated by light-initiated reactions. Among AOPs, photocatalysis has attracted the interest of researchers because it represents an effective and sustainable technology that can help solve environmental management problems, particularly pollutants in wastewater [1,2]. In the photocatalytic process, a chemical reaction is activated or its rate is changed when a semiconductor photocatalyst is irradiated by light with an energy that matches or exceeds the band gap energy of the semiconductor, resulting in excited electron-hole (e − -h + ) pairs [3]. The electrons are then promoted from the valence band (VB) to the conduction band (CB), while the holes remain in the VB. The electrons or holes interact with pollutants in the water, forming reaction intermediates. If the intermediate compounds are harmful, pollutants by removing surface-trapped electrons, thereby lowering the electron-hole recombination rate and increasing the efficiency of hole utilization for reactions such as OH − + h + → •OH [20].

Microstructural Characterization
The structural characterization of the as-prepared photocatalysts confirms that all the powders used in this study are single phases except for trace amounts of PdO in the LFP05 sample. All the compounds crystallized in a perovskite structure with an orthorhombic cell (space group Pnma) with lattice parameters close to those of LF (a = 5.5680(2) Å, b = 7.8561(3) Å, c = 5.5537(2) Å). X-ray diffraction patterns of the photocatalyst powders are shown in Figures 1 and 2. Figure 1A reports the diffraction patterns of LF, LFM05, LFM10, and LFM20; as the Mg-doping level increases, peaks broaden considerably, simultaneously shifting the Bragg angle towards a lower angle. The cell size slightly increases with increasing amounts of Mg 2+ in agreement with the ionic size of the dopant (Mg 2+ (VI) 0.72 Å vs Fe 3+ (VI) 0.645 Å). The obtained results are in agreement with data from the literature on these system [21]. presence of H2O2. The addition of H2O2 increases the photodegradation rate of organic pollutants by removing surface-trapped electrons, thereby lowering the electron-hole recombination rate and increasing the efficiency of hole utilization for reactions such as OH − + h + → •OH [20].

Microstructural Characterization
The structural characterization of the as-prepared photocatalysts confirms that all the powders used in this study are single phases except for trace amounts of PdO in the LFP05 sample. All the compounds crystallized in a perovskite structure with an orthorhombic cell (space group Pnma) with lattice parameters close to those of LF (a = 5.5680(2) Å, b = 7.8561(3) Å, c = 5.5537(2) Å). X-ray diffraction patterns of the photocatalyst powders are shown in Figures 1 and 2. Figure 1A reports the diffraction patterns of LF, LFM05, LFM10, and LFM20; as the Mg-doping level increases, peaks broaden considerably, simultaneously shifting the Bragg angle towards a lower angle. The cell size slightly increases with increasing amounts of Mg 2+ in agreement with the ionic size of the dopant (Mg 2+ (VI) 0.72 Å vs Fe 3+ (VI) 0.645 Å). The obtained results are in agreement with data from the literature on these system [21]. In Figure 1B, the diffraction patterns of LFC10 and LFG10 compared to the reference LF are reported. In LFC10, the larger ionic radius of Cu 2+ (VI) = 0.73 Å compared to Fe 3+ (VI) counterbalanced the unit cell contraction due to (i) the presence of oxygen vacancies and (ii) redox reactions in the Fe sites (the ionic radius of Fe 4+ (VI) = 0.585 Å) [22]. For LFG10, the shift toward a higher angle indicates a slight decrement of the lattice parameters in agreement with [23].
A shift in the positions of the peaks for LYF10 and LYF20, leading to an overall small reduction in cell volume, can be seen in the enlargement of Figure 2A. The substitution of the La 3+ ion (1.16 Å) with smaller Y 3+ (1.019 Å) induced an increase in the octahedral distortion (compression), which led to a reduction in the lattice parameters and unit cell volume, as previously reported [24]. In Figure 2B, LFP03 and LFP05 are reported: the peaks are slightly shifted towards low angles in the diffractograms, corresponding to their cell size increasing with increasing amounts of Pd 2+ . The ionic size of the dopant Pd 2+ (VI) was 0.86 Å, while that of Fe 3+ (VI) was 0.645 Å. Palladium oxide (PdO) was detected in the pattern of LFP05, possibly as a result of the small solubility limit of Pd in LaFeO3 [25]. However, traces of PdO cannot be excluded in LFP03 if below the detection limit. , and LFY20 are shown: the peaks are slightly shifted towards high angles, corresponding to cell size shrinking and increasing the amount of Y 3+ ; (B) X-ray diffraction patterns of LF, LFP03, and LFP05. On the right are enlargements of the (121) peak.

Brunauer-Emmett-Teller (BET) Specific Surface Area (SSA)
The specific surface area (SSA) and the crystallite size of the samples are listed in Table 1. With respect to the composition of the reference LF, which shows an SSA of 16 m 2 g −1 , the surface areas of LFM05, LFM10, LFM20, and LSF20 were enhanced, reaching a value ~20 m 2 g −1 for LFM20. The crystallite sizes calculated from the XRD analysis ranged from 18 nm (LFM20) to 45 nm (LFG10).

Sample
Nominal Composition BET (m 2 g −1 ) Crystallite Size (nm) LFC10 LaFe0.90Cu0.10O3 12 27 Figure 2. (A) X-ray diffraction patterns of LF, LFY10, and LFY20 are shown: the peaks are slightly shifted towards high angles, corresponding to cell size shrinking and increasing the amount of Y 3+ ; (B) X-ray diffraction patterns of LF, LFP03, and LFP05. On the right are enlargements of the (121) peak.
In Figure 1B, the diffraction patterns of LFC10 and LFG10 compared to the reference LF are reported. In LFC10, the larger ionic radius of Cu 2+ (VI) = 0.73 Å compared to Fe 3+ (VI) counterbalanced the unit cell contraction due to (i) the presence of oxygen vacancies and (ii) redox reactions in the Fe sites (the ionic radius of Fe 4+ (VI) = 0.585 Å) [22]. For LFG10, the shift toward a higher angle indicates a slight decrement of the lattice parameters in agreement with [23].
A shift in the positions of the peaks for LYF10 and LYF20, leading to an overall small reduction in cell volume, can be seen in the enlargement of Figure 2A. The substitution of the La 3+ ion (1.16 Å) with smaller Y 3+ (1.019 Å) induced an increase in the octahedral distortion (compression), which led to a reduction in the lattice parameters and unit cell volume, as previously reported [24]. In Figure 2B, LFP03 and LFP05 are reported: the peaks are slightly shifted towards low angles in the diffractograms, corresponding to their cell size increasing with increasing amounts of Pd 2+ . The ionic size of the dopant Pd 2+ (VI) was 0.86 Å, while that of Fe 3+ (VI) was 0.645 Å. Palladium oxide (PdO) was detected in the pattern of LFP05, possibly as a result of the small solubility limit of Pd in LaFeO 3 [25]. However, traces of PdO cannot be excluded in LFP03 if below the detection limit.

Brunauer-Emmett-Teller (BET) Specific Surface Area (SSA)
The specific surface area (SSA) and the crystallite size of the samples are listed in Table 1. With respect to the composition of the reference LF, which shows an SSA of 16 m 2 g −1 , the surface areas of LFM05, LFM10, LFM20, and LSF20 were enhanced, reaching a value~20 m 2 g −1 for LFM20. The crystallite sizes calculated from the XRD analysis ranged from 18 nm (LFM20) to 45 nm (LFG10).

Scanning Electron Microscopy (SEM) and Energy Dispersive X-ray Analysis (EDX)
The SEM micrographs shown in Figures 3 and 4 are useful for studying the morphology of the investigated samples. In particular, Figure 3 shows images of the LFC10 and LFG10 samples and a micrograph of LFM20, chosen as representative of the three samples containing magnesium. For each sample, two different magnifications (50,000× and 200,000×) are reported. On the other hand, in Figure 4, micrographs of the samples LFP05 and LFY20 (chosen as representative of the samples of their respective series) and those of the LFS20 sample are reported at two different magnifications (50,000× and 200,000×). The morphologies of all the samples studied indicate that, in general, they comprised an agglomerate of particles whose sizes ranged from ca. 20 nm to ca. 100 nm depending on the catalyst. In addition, in all cases, the particles were linked together to form corrugated sheets that were often curved and intertwined, giving rise to the formation of macropores. It is interesting to note that the morphology of the reference LF's composition, images not reported for the sake of brevity, was similar to that of the substituted LF. By analyzing the various samples in more detail, it can be observed that those that had particles of a smaller size also had a higher specific surface area. In particular, the sample LFM20, which showed the highest SSA (20 m 2 g −1 ), was the catalyst with the smallest particle size (its average size being in the range of 20-30 nm). On the contrary, the sample LFP05, with a particle size up 100 nm, showed the smallest SSA. size also had a higher specific surface area. In particular, the sample LFM20, which showed the highest SSA (20 m 2 g −1 ), was the catalyst with the smallest particle size (its average size being in the range of 20-30 nm). On the contrary, the sample LFP05, with a particle size up 100 nm, showed the smallest SSA.   Table 2 reports the percentage of metal content in all of the samples, measured using EDX analysis, compared with that of their nominal compositions. As can be observed in the table, the metal content measured using EDX analysis was generally very close to the nominal one. However, in the case of the LFM20 sample, the amount of magnesium was ca. double with respect to the nominal one, indicating an Mg-rich phase on the surface of the sample, probably due to the high amount of this element in the sample. size also had a higher specific surface area. In particular, the sample LFM20, which showed the highest SSA (20 m 2 g −1 ), was the catalyst with the smallest particle size (its average size being in the range of 20-30 nm). On the contrary, the sample LFP05, with a particle size up 100 nm, showed the smallest SSA.   Table 2 reports the percentage of metal content in all of the samples, measured using EDX analysis, compared with that of their nominal compositions. As can be observed in the table, the metal content measured using EDX analysis was generally very close to the nominal one. However, in the case of the LFM20 sample, the amount of magnesium was ca. double with respect to the nominal one, indicating an Mg-rich phase on the surface of the sample, probably due to the high amount of this element in the sample.  Table 2 reports the percentage of metal content in all of the samples, measured using EDX analysis, compared with that of their nominal compositions. As can be observed in the table, the metal content measured using EDX analysis was generally very close to the nominal one. However, in the case of the LFM20 sample, the amount of magnesium was ca. double with respect to the nominal one, indicating an Mg-rich phase on the surface of the sample, probably due to the high amount of this element in the sample.

Photocatalytic Degradation of CP and OTC
The highly performant photocatalysts on OTC degradation using UV or visible light are listed in Table S1 in Supplementary Materials. Past experimental studies have been generally performed with OTC concentrations in the range 5-50 mg L −1 , much larger than the one used in this study (0.5 mg L −1 ). Specifically, here, the concentration of the pollutant was chosen taking into account two conditions: (i) the concentration of pollutant measured in surface water is typically <1 µg L −1 in different areas [26] and (ii) this concentration must be sufficiently high for spectroscopic detection.
The ability for LF, LFY10, LFC10, and LFM10 to photodegrade CP in aqueous solutions at (i) their natural pH (pH = 6.4) and (ii) in phosphate buffered solutions (pH = 5.0) have been studied. Interestingly, it has been found that the presence of phosphate shifts the maximum absorption peak from λ = 270 nm to λ = 275 nm and decreases the absorption of CP into photocatalysts. Generally, this is ascribed to the chemical characteristics of the antibiotics and their different capabilities for forming chemical complexes. Phosphate absorption can significantly increase the number of negative charges on the photocatalyst surface, causing attraction or repulsion between phosphate and pharmaceuticals, and adsorption-site competition effects can happen due to the smaller molecular size of phosphate ions. The outcomes of our analyses on the degradation of CP are given in Table 3. C 0 and C t are the concentrations of CP before and after irradiation, respectively. Notably, only 41-22% of CP was found at a natural pH in the presence of the four photocatalysts after 240 min of visible light irradiation, whilst 72-46% of the initial CP was observed after the same irradiation time in the presence of the phosphate buffer. These results suggest that it is important to quantitatively compare the photocatalytic activities of doped-LF using an unbuffered solution for CP. Table 3. Photocatalytic degradation results reported as residual percentage of CP (calculated as C t /C 0 ·100) after 240 min of visible light irradiation in unbuffered solution of pollutant (C 0 = 5 × 10 −6 M, pH = 6.4) and in phosphate buffered solution (pH = 5.0). The photolytic degradation of OTC and CP in neat water are presented in Figure 5A,B (data named "blank"). A number of previous studies have shown that CP is susceptible to direct photochemical transformation from exposure to ultraviolet (UV-A) light [27]. CP photolytically degraded better than OTC, and the same result was found in presence of H 2 O 2 . Doped-LF-mediated heterogeneous photocatalysis was faster than pure photolysis for both molecules. Previously, it was observed that a small H2O2 addition is advantageous for the photo-oxidation of CP in the presence of LF [6]. The radical intermediate •OH formed from this oxidant from reactions with the photogenerated electrons can act as an electron scavenger, thus inhibiting the recombination of e − /h + pairs at the semiconductor surface [28] according to the following equation:

Solution
where eCB − indicates an electron excited to the conduction band.
OTC and CP showed different responses to doped-LF photocatalysts. The most extensive photodegradation of OTC, 78%, was detected with LFC10, and there was also a good response in the presence of the LFM10 photocatalyst. LSF20 showed the lowest degradation value. The most significant outcomes for CP were observed for LFM10, LFY10, and LFY20, with percentages of degradation equal to 78%, 70%, and 71%, respectively. The worst values were found with LSF20, LFG10, and LFM20. Among the doped catalysts, LSF20 showed the worst performance in both CP and OTC degradation. It seems that doping with Sr cancelled the activity of the catalyst; in fact, its activity was similar to that of the test carried out with H2O2 alone.
To compare the photocatalytic activities of LFM10 and LFC10, the reaction rate constants (k) were calculated using the pseudo first-order model (ln(Ct/C0) versus time) typically used to describe photocatalytic degradation assuming a low initial concentration of the pollutant ( Figure S2). As shown in Table 4, the apparent rate constants of OTC were determined to be 0.0051 and 0.0068 min −1 for LFM10 and LFC10, respectively, and those of CP were 0.0069 and 0.0042 min −1 for LFM10 and LFC10, respectively. Most of the removal percentage of the data in Table S1 are not comparable with ours because UV or solar radiation was used as light source. Few of these studies have been carried out using only radiation in the visible range (entries 3, 7, 8, and 9 in Table S1). Entries 3 and 7 show a very high removal efficiency (and rate constant values greater than those of solar or UV radiation) because they describe studies on composite photocatalysts, in which the enhancement of the photocatalytic performance is related to the presence of the graphene phase that causes a decrement of the recombination of photogenerated electron-hole pairs. Moreover, the unbonded π electrons of graphene provide a large absorption of OTC molecules via π-π interactions.  Doped-LF-mediated heterogeneous photocatalysis was faster than pure photolysis for both molecules. Previously, it was observed that a small H 2 O 2 addition is advantageous for the photo-oxidation of CP in the presence of LF [6]. The radical intermediate •OH formed from this oxidant from reactions with the photogenerated electrons can act as an electron scavenger, thus inhibiting the recombination of e − /h + pairs at the semiconductor surface [28] according to the following equation: where e CB − indicates an electron excited to the conduction band. OTC and CP showed different responses to doped-LF photocatalysts. The most extensive photodegradation of OTC, 78%, was detected with LFC10, and there was also a good response in the presence of the LFM10 photocatalyst. LSF20 showed the lowest degradation value. The most significant outcomes for CP were observed for LFM10, LFY10, and LFY20, with percentages of degradation equal to 78%, 70%, and 71%, respectively. The worst values were found with LSF20, LFG10, and LFM20. Among the doped catalysts, LSF20 showed the worst performance in both CP and OTC degradation. It seems that doping with Sr cancelled the activity of the catalyst; in fact, its activity was similar to that of the test carried out with H 2 O 2 alone.
To compare the photocatalytic activities of LFM10 and LFC10, the reaction rate constants (k) were calculated using the pseudo first-order model (ln(C t /C 0 ) versus time) typically used to describe photocatalytic degradation assuming a low initial concentration of the pollutant ( Figure S2). As shown in Table 4, the apparent rate constants of OTC were determined to be 0.0051 and 0.0068 min −1 for LFM10 and LFC10, respectively, and those of CP were 0.0069 and 0.0042 min −1 for LFM10 and LFC10, respectively. Most of the removal percentage of the data in Table S1 are not comparable with ours because UV or solar radiation was used as light source. Few of these studies have been carried out using only radiation in the visible range (entries 3, 7, 8, and 9 in Table S1). Entries 3 and 7 show a very high removal efficiency (and rate constant values greater than those of solar or UV radiation) because they describe studies on composite photocatalysts, in which the enhancement of the photocatalytic performance is related to the presence of the graphene phase that causes a decrement of the recombination of photogenerated electron-hole pairs. Moreover, the unbonded π electrons of graphene provide a large absorption of OTC molecules via π-π interactions.

Photocatalytic Degradation of CP and OTC
Generally, the preliminary adsorption of substrate molecules on the surface of a catalyst is necessary for highly efficient photocatalytic degradation [29]. Larger surface areas provide active sites for the adsorption of reagent molecules. The adsorption of molecules on a metal-oxide surface is influenced by the acid-base properties of the surface. Some authors have reported the point of zero charge (PZC) for LF and related oxides. The PVC is a pH of 8.9 for LF [7] [32], suggesting that the surface charge of catalysts is positive when pH < 6.2 as in the case of our experiments. OTC exists predominantly as a cation at pH < 3.6 when the dimethylammonium group is protonated, as a zwitterion between pH 3.6 and 7.5 (resulting from the loss of proton from the phenolic diketone moiety), and as an anion at pH > 7.5 (resulting from the loss of protons from the tricarbonyl system and phenolic diketone moiety) [33]. In this study, the OTC solution was buffered at pH = 5.0, so OTC has zwitterionic form (see Figure S3). Figure 6 shows OTC degradation as a function of the SSA of the photocatalysts (A), and their calculated crystallite size (B). Two catalysts are missing because of the following reasons: (i) LSF20 does not show significant photocatalytic activity ( Figure 5A) and (ii) LFP05 is excluded due to the presence of PdO nanoparticles detected from the XRD analysis. In both graphs, the points lay roughly on a straight line, except for the LFC10 photocatalyst. In yellow is the 95% confidence interval for the linear interpolation (in red) of the points. The variation in OTC degradation for doped-LF photocatalysts is most likely the result of an SSA-dependent adsorption on the catalyst surface of the OTC molecules. This relation between the SSA of the photocatalyst and the photocatalytic degradation of OTC indicates that surface reactions are predominant compared to radical reactions in the solution. However, the SSA is not sufficient to explain all results, since the SSA of LFC10 is smaller than, for example, that of LF. Previously, photocatalyst stability was assessed using leaching experiments under solar light in the absence of a pollutant [34]. No significant amounts of Fe, Cu, or La were measured with respect to the lowest limits of their quantification values (Fe = 0.05 mg/L, Cu = 0.03 mg/L and La = 0.1 mg/L). For this reason, a contribution via Cu 2+ complexation in the solution is excluded. A possible explanation for the better performance of LFC10 could be the presence of oxygen vacancies, as reported in Cu-doped LaAlO 3 , which are favorable for the dissociation of H 2 O 2 and the generation hydroxyl radicals [35]. As expected, the crystallite size dependence of OTC degradation shows a similar behavior to SSA.

BET Specific Surface Area (SSA) and CP Degradation
CP possesses a carboxylic acid group (pK a1 = 6.1) and an amine group in the piperazine moiety (pK a2 = 8.7) [36]. It can exist predominantly as a cation at pH < 6.1, as a zwitterion between pH 6.1 and 8.7, and as an anion at pH > 8.7. Surface complexation with positively charged sorbents can occur with deprotonated carboxylate and keto groups. Figure 7 shows CP degradation as a function of the SSA of the photocatalysts and their calculated crystallite size. Unlike what is observed with OTC, the results suggest that microstructural features have poor influence on the extent of the degradation. In this study, the initial pH of the solution was about 6.4, so CP zwitterionic and cationic forms were predominant. During the degradation reactions, the pH dropped just below 6.1 due to the formation of inorganic acids, such as HF and HNO 3 , and low molecular weight organic species, such as carboxylic acids [37]. In general, pH affected the adsorption of the pollutant on the catalyst. When the solution pH was lower than 6.1, the surface of the doped-LF oxides was positively charged, and the catalyst exhibited electrical repulsion that hindered the adsorption of CP cations; thus, the reaction efficiency dropped. This fact is evident from an analysis of the results obtained from the photocatalytic tests performed with CP at a pH of 5 (see Table 3). The degradation of CP observed at a pH of 5 indicates that the reaction occurred only in the homogeneous phase and, furthermore, that the presence of the catalyst negatively affected the degradation of CP as a result of a light shielding effect. In fact, the degradation rate of CP in the presence of a photocatalyst was always lower than that of CP in the presence of H 2 O 2 alone. On the contrary, the tests carried out at an initial pH of 6.4 indicate that the degradation of CP in the presence of a photocatalyst was generally slightly higher than that of CP in the presence of H 2 O 2 alone. This indicates that the homogeneous reaction is the prevailing one and, therefore, at this pH, a leveling in the amount of CP degraded is observed.

BET Specific Surface Area (SSA) and CP Degradation
CP possesses a carboxylic acid group (pKa1 = 6.1) and an amine group in the piperazine moiety (pKa2 = 8.7) [36]. It can exist predominantly as a cation at pH < 6.1, as a zwitterion between pH 6.1 and 8.7, and as an anion at pH > 8.7. Surface complexation with positively charged sorbents can occur with deprotonated carboxylate and keto groups. Figure 7 shows CP degradation as a function of the SSA of the photocatalysts and their calculated crystallite size. Unlike what is observed with OTC, the results suggest that microstructural features have poor influence on the extent of the degradation. In this study, the initial pH of the solution was about 6.4, so CP zwitterionic and cationic forms were predominant. During the degradation reactions, the pH dropped just below 6.1 due to the formation of inorganic acids, such as HF and HNO3, and low molecular weight organic species, such as carboxylic acids [37]. In general, pH affected the adsorption of the pollutant on the catalyst. When the solution pH was lower than 6.1, the surface of the doped-LF oxides was positively charged, and the catalyst exhibited electrical repulsion that hindered the adsorption of CP cations; thus, the reaction efficiency dropped. This fact is evident from an analysis of the results obtained from the photocatalytic tests performed with CP at a pH of 5 (see Table 3). The degradation of CP observed at a pH of 5 indicates that the reaction occurred only in the homogeneous phase and, furthermore, that the presence of the catalyst negatively affected the degradation of CP as a result of a light shielding effect. In fact, the degradation rate of CP in the presence of a photocatalyst was always lower than that of CP in the presence of H2O2 alone. On the contrary, the tests carried out at an initial pH of 6.4 indicate that the degradation of CP in the presence of a photocatalyst was generally slightly higher than that of CP in the presence of H2O2 alone. This indicates that the homogeneous reaction is the prevailing one and, therefore, at this pH, a leveling

Microstructural Characterization
The powder X-ray diffraction patterns of the catalysts were recorded using a Bruker D8-Advance powder diffractometer equipped with a Cu kα X-ray source and a Lynxeye XE-T ® solid-state detector. The patterns were recorded in an interval of 10-90 • 2θ with a step of 0.01 • and a counting time of 1 s per step. X-ray data were used to calculate domain size using the Scherrer equation. Brunauer-Emmett-Teller (BET) specific surface area (SSA) determination was performed with nitrogen absorption on about 500 mg of the samples using a Micrometric Tristar 3000 automated gas-adsorption analyzer.

Scanning Electron Microscopy (SEM) and Energy Dispersive X-ray Analysis (EDX)
Scanning electron microscopy (SEM) was performed using an FEI Quanta 200 ESEM microscope, operating at 20 kV on specimens from which a thin layer of gold had evaporated. On the other hand, an electron microprobe used in an energy dispersive mode (EDX) was employed to obtain information on the actual metal-content ratio present in the samples.

Photocatalytic Studies
Photocatalytic degradation reactions were carried out using a Ryonet reactor equipped with 6 fluorescent lamps (daylight, 8W, GE lighting 10055-F8T5/D) emitting in the 380-780 nm region. The temperature was kept constant at 28 ± 1 • C through a liquid cooling system. In the typical process, 2.6 mg of photocatalyst powder was added to 20 mL of a 5.0 × 10 −6 M aqueous solution of CP or OTC with the presence of 10 −2 M H 2 O 2 . The mixture was stirred in the dark for 20 min in a Pyrex glass tube in order to allow for an adsorption/desorption equilibrium on the catalyst surface. Then, the 6 lamps were turned on for 4 h at different time intervals (t = 0, 30, 60, 120, and 240 min), and aliquots of the reacting suspension (2.5 mL) were taken. The samples were centrifugated for 5 min at 350 rpm (Scharlab BL-8), and their supernatants were analyzed on the spectrophotometer (see Section 2.5). The photocatalytic activities of the samples were evaluated by monitoring the degradation of CP in a buffered solution (buffer phosphate, 100 mM pH = 5.0) and in an unbuffered CP solution (initial solution pH = 6.0, and about 6.4 when the photocatalysts were also present). The degradation of OTC was evaluated only in the buffered solution (buffer phosphate, 100 mM pH = 5.0) since, at pH 5.0, OTC cannot be photolyzed under visible light because of its poor visible light absorption [38]. All degradation tests were repeated twice.

UV-Vis Spectroscopy
The absorption spectra were measured using an ultraviolet-visible (UV-Vis) doublebeam spectrophotometer (Jasco V-650) with a 10-mm light path and quartz cuvettes. Full spectra were taken in order to monitor any spectral change that may have occurred. The degradation of CP and OTC were calculated using the formula C t /C 0 , where C 0 and C t are the concentrations of the pollutant in the solution before and after irradiation, respectively, at a set time (t). Degradation values are the average of two independent assays. The main absorption peaks were detected at 270 nm for CP and 350 nm for OTC. Figure 8 shows the absorption spectra of the investigated molecules.

UV-Vis Spectroscopy
The absorption spectra were measured using an ultraviolet-visible (UV-Vis) doublebeam spectrophotometer (Jasco V-650) with a 10-mm light path and quartz cuvettes. Full spectra were taken in order to monitor any spectral change that may have occurred. The degradation of CP and OTC were calculated using the formula Ct/C0, where C0 and Ct are the concentrations of the pollutant in the solution before and after irradiation, respectively, at a set time (t). Degradation values are the average of two independent assays. The main absorption peaks were detected at 270 nm for CP and 350 nm for OTC. Figure 8 shows the absorption spectra of the investigated molecules.

Conclusions
Many studies focusing on heterogeneous photocatalysis for water treatment have reported on the synthesis of novel semiconductor oxides, their physico-chemical characterizations, and the degradation of model compounds. We have shown herein that the selection of the substrate (model compound) is critical. To obtain reliable conclusions, it is good to use one (or more) model molecules exhibiting electrostatic attraction with the surface of the photocatalyst and also one exhibiting electrostatic repulsion.
In this study, pure and doped semiconductor oxides (La1-xAxFeO3 A = Y; Sr and LaFe1-xBxO3 B = Cu, Ga, Mg, Pd) were prepared using the sol-gel method and used for the photocatalytic degradation of model pollutants, the OTC and CP antibiotics in water. LFM10 and LFC10 are able to remove 71% and 78% of OTC (C0 = 5·× 10 −6 M, buffer pH = 5.0) in 240 min in the presence of H2O2 and under visible light irradiation, respectively. The specific surface area (SSA) and doping type are the main factors affecting degradation capacity. LFM10, LFY10, and LFY20 photocatalysts showed a remarkable photocatalytic activity degrading CP (78%, 71%, and 70% of CP removal in 240 min, respectively) using starting conditions C0 = 5·× 10 −6 M and a natural pH of 6.4. OTC and CP exist predominantly as a cation at pH < 3.6 and pH < 6.1, respectively. As a consequence, unlike what is observed with OTC, when the electrostatic repulsion between the pollutant (CP) and the oxide surface is predominant (pH below 6.1), the microstructural features have poor influence on the extent of degradation.

Conclusions
Many studies focusing on heterogeneous photocatalysis for water treatment have reported on the synthesis of novel semiconductor oxides, their physico-chemical characterizations, and the degradation of model compounds. We have shown herein that the selection of the substrate (model compound) is critical. To obtain reliable conclusions, it is good to use one (or more) model molecules exhibiting electrostatic attraction with the surface of the photocatalyst and also one exhibiting electrostatic repulsion.
In this study, pure and doped semiconductor oxides (La 1-x A x FeO 3 A = Y; Sr and LaFe 1-x B x O 3 B = Cu, Ga, Mg, Pd) were prepared using the sol-gel method and used for the photocatalytic degradation of model pollutants, the OTC and CP antibiotics in water. LFM10 and LFC10 are able to remove 71% and 78% of OTC (C 0 = 5 × 10 −6 M, buffer pH = 5.0) in 240 min in the presence of H 2 O 2 and under visible light irradiation, respectively. The specific surface area (SSA) and doping type are the main factors affecting degradation capacity.
LFM10, LFY10, and LFY20 photocatalysts showed a remarkable photocatalytic activity degrading CP (78%, 71%, and 70% of CP removal in 240 min, respectively) using starting conditions C 0 = 5 × 10 −6 M and a natural pH of 6.4. OTC and CP exist predominantly as a cation at pH < 3.6 and pH < 6.1, respectively. As a consequence, unlike what is observed with OTC, when the electrostatic repulsion between the pollutant (CP) and the oxide surface is predominant (pH below 6.1), the microstructural features have poor influence on the extent of degradation.

Conflicts of Interest:
The authors declare no conflict of interest.